Impact of Groundwater Quality Status on its Sustainable Use Case study: Northwest of ,

Samir R. Awad, Zeinab M. El Fakharany

Associate Professor, Research Institute for Groundwater (RIGW), National Water Research Center (NWRC) Email: [email protected], ORCID iD: https://orcid.org/0000-0001-8251-8492

Abstract: The research area is located in the northwest of Giza city. The main objective of the study is to evaluate the groundwater quality status and the hazardous impacts for sustainable uses. Chemical results showed that the total dissolved solids (TDS) in drains are ranging between 633 mg/l and 1746 mg/l and nitrate (NO3) concentrations range from 48 mg/l to 88 mg/l. High TDS in the groundwater reaching 4768 mg/l and high concentrations of nitrate more than 45 mg/l are found only in the western and southwestern parts of the study area referring to agricultural and domestic wastes. Simulation of groundwater flow using MODFLOW indicated that the aquifer in the modeled area is recharged dominantly from excess irrigation water and leakage from irrigation network. Both MODPATH and MT3DMS results confirmed that contaminants migrate downward and extending into the unconfined highly vulnerable aquifer part, which affected the groundwater sustainable use. [Samir R. Awad, Zeinab M. El Fakharany. Impact of Groundwater Quality Status on its Sustainable Use Case study: Northwest of Giza, Egypt. Nat Sci 2020;18(1):155-170]. ISSN 1545-0740 (print); ISSN 2375-7167 (online). http://www.sciencepub.net/nature. 21. doi:10.7537/marsnsj180120.21.

Keywords: Groundwater; quality; wastewater; MODFLOW; sustainable use; Giza, Egypt

1. Introduction and human activities on groundwater and related Greater is the most populous area in Egypt environment (Namitha et al. 2019, Zhou and Li, 2011, with estimates of around 18 million citizens. The Loucks et al., 1985). Moreover, groundwater modeling domestic wastewater quantity raised due to high gained wide application due to the availability of intensity of the population. There are approximately modern software packages and powerful computers. 164 wastewater treatment plants in Egypt mainly Many studies have been followed out on numerical execute the secondary treatment. Only three plants groundwater modeling for assessment and execute primary treatment: two in and one management (Namitha et al. 2019, Khalaf and Gad, in Cairo (Abu Rawash wastewater treatment plant 2015, Chao et al. 2010, Senthilkumar and Elango, WWTP). The capability of the current primary Abu 2004, Balazova et al. 2002), as well as studies deal Rawash WWTP in Cairo is 1.2 million m3/day, which with the pollution and the contamination of does not meet the legal requirements. Excess sewage groundwater (Zeidan et al., 2013, El-Araby,2008, amounts are discharged without treatment causing Shamrukh,2001). Therefore, the present study aims at water pollution in drains and subsequently evaluating the groundwater quality status in the contributing pollution loads to the branch. northwest of Giza city and the hazardous impacts for Only primary treatment will remain insufficient to sustainable use. satisfy environmental and legal limitations. the The research area is present in the northwest of provision of at least secondary treatment facilities is Giza city among longitudes from 31° to 31° 10' E and essential to meet the conditions and to improve the latitudes from 30° to 30° 10' N (Figure 1). There is a water quality and environment of the receiving water main wastewater treatment plant at Abu Rawash area bodies. The wastewater utilities were created in 1981 with maximum effluents 1,450,000 m3/day and 1979 by Presidential Decrees (MHUUD, 2010). (Mohamed, 2015). The whole drainage system In Egypt, groundwater is performing a vital role discharges treated with untreated wastewater into in development. Therefore, it is necessary to take in Barakat drain that reaches the extension of El Mouhit mind the hydrogeology of the groundwater aquifer and drain and then El Rahawy drain that discharges finally its vulnerability to pollution to protect it from huge amounts of wastewater at the Rosetta branch, pollution. Nowadays, groundwater model has become therefore it has harmful impacts on its water quality an essential tool for hydrogeologists to perform due to its high organic loads (Mohamed, 2015). various tasks including helps in formulating the management strategy, the assessment and forecast of 2. Description of the Study Area groundwater, the discovery of groundwater pollution The present study area is marked by a gentle

155 Nature and Science 2020;18(1) http://www.sciencepub.net/nature NSJ slope in topographic features, where ground elevation  Old alluvial plain covers the western part varies between less than 20 m +msl at the east and forming gravel terraces (Said, 1990). It contains new greater than 50 m + msl at the southwestern portions reclaimed lands irrigated using groundwater and partly (EGSA, 1997). The geomorphologic features in the reused drainage water to cover water the shortage in study area include i) The young alluvial plain; ii) The some locations. old alluvial plain, and iii) El Hassana dome and  El Hassana dome is a geologic structure bounding slopes. covering an area of one square kilometer, which is  Young alluvial plains cover the eastern part located about 23 km northwest from Cairo (Said, that contains the old cultivated lands, irrigation canals, 1990). drains and towns with the extensive population.

Figure 1: Location of the present study area on Google earth image.

The air temperature (T) rises in summer with semi-pervious layers (Figure 2). There is a direct maximum average values exceeding 40 ºC during contact between surface water and subsurface. There July, while minimum average values below 14are are many open drains in the study area that are giving measured during January. The relative humidity (R.H.) a chance for the wastewater and excess irrigation reaches its maximum average values of 55% in July water to move down to the subsurface causing and August and its minimum values of 37% in April recharge to the groundwater aquifer. (Sharaky et al. 2017). Evaporation intensity (Ev) is a The geological map, as shown in figure 2, shows significant factor affecting water quality, particularly the surface outcrops of different geological formations where groundwater is close to the ground surface. The and structures in the study area (EGPCO, CONOCO, rainfall effect on the surface and groundwater is 1987, RIGW, 1989). The Quaternary aquifer consists insignificant, especially during summer due to limited of consecutive layers of sand and gravels intercalated quantity (UNDP, 2013). by clay lenses. Its maximum thickness is about 200 m in the northern part and decreases to the south 3. Hydrogeological Setting reaching 100 m in the south. Also, the aquifer The surface water system includes the El thickness vanishes westward until the Quaternary Mansuriya canal that is passing through pervious and sediments overlap with the tertiary sediments of

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Miocene, Oligocene or older rocks (Figure 3). The saturated with groundwater especially northeastern thickness of Miocene sediments is about 50 m of sand portion. The groundwater exists dominantly under free and clay. Oligocene basalts are occasionally water table conditions (unconfined) to semi-confined underlying the Miocene and overlying the Oligocene where semi-pervious clay cap covers the aquifer, sediments. The layer forming the Quaternary aquifer is especially in the eastern parts.

Figure 2: Geological map of the study area (after EGPCO, CONOCO, 1987).

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Figure 3: Hydrogeological cross sections (after RIGW, 1989).

Table 1: locations and sources of water samples. Sample Code Well Depth (m. -GL) Depth to Water Table (m. -GL) Groundwater Levels (m. +msl) W1 65 6,5 12 W2 48 7.3 11.5 W3 62 11.5 12.6 W4 70 1.5 14 W5 35 8.5 12 W6 65 10 11 W7 56 5 12.5 W8 54 10.5 12 W9 35 8 12.5 Mn. C El Mansouriya Canal Dn1 El Mouhit Drain Dn2 El Mansouriya Drain Dn3 El Mouhit Drain

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4. Material and Methods spectrophotometer and the highly sensitive analytical Geological, hydrogeological and hydrochemical methods have been used. Thirteen water samples have data have been collected and inventoried in the been examined for dissolved chemical constituents fieldwork and used for the present study (Table 1). (EC, pH, K, Ca, Na, Mg, HCO3, SO4, Cl, NO3 and Data about groundwater levels were collected and some trace elements. measured in wells to update the groundwater levels The sodium adsorption ratio (SAR) is a simple map. Then, groundwater vulnerability map used for method used to evaluate the danger of high sodium quantifying the availability of pollutants from concentrations in irrigation water (Freeze and Cherry, hazardous sources to reach groundwater. 1979). Wilcox classification diagram has used to Standard methods of water sampling and distinguish the groundwater samples for irrigation uses chemical investigations was applied for major cations (Wilcox 1955). Electrical conductivity (EC) shows the and anions, nutrients and trace elements contents in salinity hazard and SAR ratio shows the alkalinity groundwater and surface water samples. All these hazard. Water types divided into four categories (S1, chemical analyses have been carried out in the Central S2, S3, S4) based on salinity hazard and another four Laboratory, NWRC according to the standard methods categories (C1, C2, C3, C4) based on sodium hazard (APHA, 2017). Methods of chemical titration by as shown in table 2 (Wilcox, 1955). standard indicators; flame photometer;

Table 2: Classification of Water Suitability for Irrigation (After Wilcox, 1955). EC (uS/cm) at 25° Salinity Na Class Class SAR Usage C content content C1 <250 Low S1 < 10 Low Can be used for all soils 10 - C2 250-750 Medium S2 Medium used for coarse texture, soils of good permeability 18 18 - Can produce harmful effects and good soil management is C3 750-2250 High S3 High 26 essential C4 >2250 Very high S4 >26 Very high Not satisfactory for irrigation purposes

The groundwater flow model software (Visual  The southern boundary is a specified head MODFLOW), based on the finite-difference technique boundary coinciding with the piezometric headlines (McDonald and Harbaugh, 1988), has been used to ranging from 12 m +msl to 13.5 m +msl. simulate the hydrogeological conditions of the The sources of the data include the RIGW groundwater aquifer system in the study. The modeled database and field measurements. Hydrogeological area extends with a width of 10.5 km and a length of studies showed a semi-confined groundwater aquifer 18 km, with an area of about 189 km2. The grid, of under the old lands to the east, while in the western rectangular shape, covered the modeled area and fringes the aquifer is phreatic due to the loss of the consisted of 361 rows and 211 columns (Figure 4). superficial clay cap layer (RIGW, 1992). The Three layers have been modeled; 1) clay cap layer horizontal hydraulic conductivity of the groundwater covering the aquifer with a thickness 15 m to the east aquifer ranges from 50 to 75 m/day and decreases to and vanishing westward (Al-Agha et al. 2015), 2) 40 m/day in the phreatic aquifer to the west of the Quaternary aquifer layer with a maximum depth of study area. The horizontal permeability of the semi 200 m, and 3) Miocene/Oligocene aquifer layer pervious clay cap layer ranges from 1.0 to 2.0 m/day, located in the southwestern part of the modeled area. while the vertical permeability ranges from 0.01 to 0.2 The boundary condition was selected depending m/day (RIGW, 2002). on the hydrogeological situation of the modeled area The particle tracking module (MODPATH) used (Figure 4). to show pollutant transport and to calculate three-  The northern boundary is a constant head dimensional particle tracking with pathlines using boundary coinciding with El Rayah El Nasseri steady-state flow simulation achieved by MODFLOW channel. (Pollock, 2017). The pathlines outline the transport  The eastern boundary is a constant head pathlines and travel time of particles due to boundary coinciding with El Mouhit drain. groundwater flow.  The western boundary is a specified head MT3DMS is a groundwater three-dimensional boundary coinciding with the piezometric head line 12 solute transport model used to simulate contaminant m +msl. transport in groundwater aquifer (Zheng and Wang,  The southwestern boundary is no flow 1999). That model has been designed to be used after boundary coinciding with the limestone plateau. the construction and calibration of the flow model

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(MODFLOW) at the beginning. Therefore, the solute processes as wastewater contaminants on the aquifer transport model (MT3DMS) was used to simulate and system. forecast the effect of TDS and NO3 transportation

Figure 4: Grid and boundary conditions.

5. Results and Discussion maps serve as guidelines for land use and the The present study revealed groundwater status in development of policies for groundwater protection the research area and its sustainability use in the (UNESCO-ACSAD, 1995). The concept of following: vulnerability has evolved in the past for the 5.1. Groundwater Level assessment of contamination risk placed upon aquifers Measured and collected data about groundwater by human activities. In the newly planned areas for levels (Table 1) used to update the groundwater levels projects as industrial, agricultural, urban…etc, Actions map (Figure 5). The depth to water table is about 1 m for groundwater protection must be taken according to in the northeastern part and increases southward to its vulnerability. The most important hydrogeological more than 7 m and westward to more than 12 m along characteristics that influence groundwater the western fringes. The groundwater level in the west vulnerability are the thickness of the covering clay is about 12 m +msl, to about 16 m +msl in the east cap; recharge rate to groundwater; and depth to the (Figure 5). The groundwater flows mainly towards the groundwater table (RIGW and IWACO, 1990, Al- west indicating aquifer recharge mainly from surface Adamat and Al-Shabeeb, 2017). Therefore, water and excess irrigation water. Groundwater vulnerability map was drawn to quantify 5.2. Groundwater vulnerability the availability of pollutants to reach groundwater Groundwater vulnerability map used for (Figure 6). The resultant vulnerability zones in the quantifying the availability of pollutants from research area are as follow: hazardous sources to reach groundwater. Vulnerability

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Figure 5: Updated groundwater levels map based on collected data (m +msl).

- Moderate vulnerability zones: These include The results of chemical analyses for groundwater parts characterized by a thin clay cap and deep samples, (Table 3), and those for surface water groundwater table. Groundwater in such areas could samples, (Table 4), have been used for drawing be polluted and some cautions must be considered distribution maps of different dissolved chemical while planning for new projects in such areas. parameters in groundwater. These maps represent the - High vulnerability zones: These areas are trends of increase or decrease of elements in present in the west where the clay cap is absent. groundwater. Evaluation of water uses for drinking are Groundwater in these areas could be easily polluted based on guidelines of World Health Organization and severe cautions must be recognized when planning (WHO, 2011) and the Egyptian Ministry of Health for developing such areas. (EMH, 2007) and the guidelines of FAO, 1985 for 5.3. Water quality assessment irrigation water.

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Figure 6: Distribution map of groundwater vulnerability zones.

Table 3: Chemical analysis for groundwater samples. Sample Code W1 W2 W3 W4 W5 W6 W7 W8 W9 Drinking Guidelines Irrigation Guidelines pH (Value) 8.18 7.83 7.93 8.9 7.75 7.64 8.05 7.59 7.91 6.5-8.5 6.5-8.5 EC (mmhos/cm) 1.755 1.51 1.234 1.418 0.96 7.45 1.1 2.41 1.13 1.6 3.1 TDS (mg/l) 1124 966 789 907 612 4768 705 1507 794 1000 2000 K+ (mg/l) 14 8 12 8 8 15 5 17 5

Na+ (mg/l) 160 190 120 155 62 1251 85 248 97 200

Mg2+ (mg/l) 51 27 37 34 38 60 33 69 63 150

Ca2+ (mg/l) 156 86 99 86 77 328 104 124 44 200

Cl- (mg/l) 170 275 122 157 85 1962 107 380 124 250 355 2- SO4 (mg/l) 287 150 157 114 140 1084 147 320 132 250 - HCO3 (mg/l) 351 200 331 395 278 390 326 350 329 520 2- CO3 (mg/l) 0 0 0 0 0 0 0 0 0 - NO3 (mg/l) 50 40 2 6 8 138 2 50 40 50 135 NO - (mg/l) 0.2 0.2 0.2 0.2 0.2 0.2 0.2 0.2 0.2 1 2 Al (mg/l) 0.006 0.005 0.006 0.006 0.005 0.006 0.006 1.564 0.28 0.2 20 Ba (mg/l) 0.034 0.287 0.066 0.099 0.612 0.023 0.073 0.101 0.7 -- Cr (mg/l) 0.001 0.042 0.001 0.001 0.027 0.001 0.001 0.05 1

Cu (mg/l) 0.011 0.081 0.013 0.01 0.075 0.015 0.012 2 5

Fe (mg/l) 0.008 0.298 0.008 0.008 3.279 0.008 0.02 0.624 0.3 20 Pb (mg/l) 0.003 0.001 0.003 0.003 0.001 0.003 0.003 1.773 0.01 10

Mn (mg/l) 0.005 0.368 0.005 0.005 1.509 0.005 0.092 0.427 0.4 10 Ni (mg/l) 0.091 0.01 0.004 0.005 0.001 0.004 0.004 1.077 0.07 2

Zn (mg/l) 0.001 0.323 0.001 0.001 0.667 0.001 0.001 5 10

T.Hard. (mg/l) 599 328 399 355 349 1065 393 500

SAR (Value) 2.84 4.56 2.61 3.58 1.44 16.66 1.86 2.20 - 10

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Table 4: Chemical analysis for surface samples. Mn. C Dn1 Dn2 Dn3 Mn. C Dn1 Dn2 Dn3 - pH (Value) 7.7 7 8.1 7.4 NO3 (mg/l) 4.3 88 80 48 EC (mmhos/cm) 0.55 2.75 1.96 0.99 Al (mg/l) 0.056 0.006 0.006 0.006 TDS (mg/l) 342 1746 1203 633 Ba (mg/l) 0.038 0.033 0.034 0.026 K+ (mg/l) 5 16 17 15 Cr (mg/l) 0.001 0.001 0.001 0.001 Na+ (mg/l) 39 513 312 122 Cu (mg/l) 0.037 0.068 0.04 0.026 Mg2+ (mg/l) 14 41 24 27 Fe (mg/l) 0.011 0.008 0.008 0.043 Ca2+ (mg/l) 37 92 81 54 Pb (mg/l) 0.003 0.003 0.003 0.003 Cl- (mg/l) 44 542 394 97 Mn (mg/l) 0.005 0.018 0.005 0.069 2- SO4 (mg/l) 35 204 147 62 Ni (mg/l) 0.004 0.006 0.001 0.006 - HCO3 (mg/l) 168 338 228 256 Zn (mg/l) 0.001 0.001 0.001 0.001 2- CO3 (mg/l) 0 0 0 0 SAR (Value) 1.82 9.76 8.84 3.05

5.3.1. Surface water assessment for domestic uses water in the area. The total dissolved salts (TDS) in El Mansuryia 5.3.2. Groundwater assessment for domestic uses canal is quite low reaching 342 mg/l, while the TDS The total dissolved salts (TDS) in the values in El Mouhit and El Mansuriya drains ranges groundwater samples ranged between 612 mg/l and between 633 mg/l and 1746 mg/l. High nitrate (NO3) 4768 mg/l. Figure 7 showed that fresh to brackish concentrations are detected in drains ranging from 48 groundwater (TDS < 1500 mg/l) dominated the area. mg/l to 88 mg/l. These high concentrations could be The high TDS (>1500 mg/l) in the south and referred to receiving considerable amounts of southwestern parts could be referred to infiltrated and agricultural and domestic wastes. The wastewater mixed domestic and industrial wastewater with treatment plant at Abu Rawash is not enough to treat dissolution and leaching of salts from the aquifer all wastewater due to huge quantities of drainage sediments.

Figure 7: Distribution map of groundwater salinity (TDS).

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The nitrate concentration in groundwater samples (Farrag et al, 2016). In the present study, trace varied from 2 mg/l to 138 mg/l (Table 3). The elements that analyzed in water samples are Al3+, groundwater is mostly dominated by low nitrate Ba2+, Cr2+, Cu2+, Fe2+, Mn2+, Ni2+, Pb2+, and Zn2+. concentrations less than 45 mg/l as shown in figure 8. Based on the limits presented by WHO (2011) and High concentrations of nitrate (> 45 mg/l) are EMH, (2007), the concentrations of all analyzed trace observed in the west and southwestern portions elements in both surface and groundwater samples are indicating pollution from domestic and agricultural within suitable limits for the different water uses. The wastewater especially in high vulnerability areas to low contents of groundwater trace elements could be pollution. referred to cation exchange and adsorption processes in the aquifer especially in locations where a thin clay Beside the major elements, some heavy metals cap is present and where carbonate material is present (trace elements) are of special and considerable through the aquifer sediments. importance for the study of groundwater quality

Figure 8: Nitrate distribution in Groundwater.

5.3.3. Groundwater assessment for irrigation permeability soils. Some samples in the southwestern The TDS values of the groundwater (Table 3 and part have medium (10-18) SAR content (Wilcox Figure 7) indicate suitable water for irrigation without classification), which indicating harmful water for any problem except in the southwestern location irrigation, which means a need for certain where TDS values of groundwater exceed 2000 ppm management techniques to prevent or decrease that (Figure 7). While the TDS of the other locations risk by adding Gypsum to the soil to increase the increased due to the impact of irrigation water and calcium to improve sodium/calcium ratio as shown in leaching of salts. The tendency of increasing the TDS the following equation. of the groundwater will be predicted by using a 2Na clay + CaSO4 Ca clay + Na2SO4 mathematical model. AQUACHEM hydrochemical software has been The values of SAR in groundwater samples used to construct the Wilcox diagram for samples of range between 1.44 and 16.66 with an average of 4.58 the present study as shown in figure 10. According to (Table 3). As shown in figure 8, most of groundwater Wilcox Diagram, most groundwater samples are found samples have low SAR content (<10) indicating in C2-S1, C3-S1 and C3-S2 classes indicating suitable suitable water for irrigation in coarse textured good water for irrigation with most crops in most soils.

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Some samples are plotted in C4-S3 class indicating Figure 5), against the calculated heads. The calibration unsuitable water for irrigation under common has been achieved through trial and error by adjusting circumstances due to very high salinity risk. the recharge rate and hydraulic conductivity until a 5.4. Numerical Model Results good match between the calculated and observed head Prior to prediction runs, the model has been values has been obtained. Figure 11 represents calibrated in the steady state conditions by comparing calculated calibrated piezometric head in the modeled the available historical data and the measured area. groundwater levels (observed heads) (Table 1 and

Figure 9: Distribution map of sodium adsorption ratio (SAR) in Figure 10: Wilcox diagram for groundwater groundwater. and surface water samples.

Figure 11: Calculated calibrated piezometric heads in the modeled area.

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Figure 12 illustrates chart for steady state water boundary, therefore the leakage to the aquifer from El balance (budget) given by MODFLOW simulation of Rayah El Nasseri and El Mansuriya canal is about the hydrogeological system in the modeled area. The 12604 m3/day and discharge out from the aquifer is MODFLOW water budget showed the following facts: about 561 m3/day.  The flow to the aquifer through boundary is  Recharge from surface activities to the about 51745 m3/day and the flow out from the aquifer aquifer is about 7985 m3/day. through boundary is about 56542 m3/day. Thus, the analysis of the water budget indicated  The extraction through pumping wells from recharging the aquifer through leakage from irrigation the study area is about 51250 m3/day and discharge by network and surface activates. Therefore, the aquifer drainage through El Mouhit drain is about 613 m3/day. in the modeled area is renewable and affected by  Canals was added to the model as a river surface activates.

Figure 12: Calculated water balance (budget) in the modeled area.

Figure 13: Calculated MODPATH results in the modeled area.

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The travel time of particles with groundwater The MT3DMS quality model has been used for flow was set to 50 years (life time for sustainable prediction of the effect of nitrate and total dissolved development). Results of MODPATH indicated that solids on the groundwater quality status. Results of the water flows and also drain pollutants transport MT3DMS model regarding TDS concentration mainly from northeast to southwest and from east to (Figures 14a, b) indicated that the groundwater salinity north at wastewater treatment plant (Figure 13). This (TDS) reaches to more than 1200 mg/l along the drain indicates recharging the aquifer in the modeled area route, then decreases to reach 400 mg/l outside at a from the surface water. Therefore, the aquifer is distance of 1 km far from the drain route. Predictions renewable and surface activities affected on it. The showed that the TDS concentration could be increased model indicated that the velocity of groundwater flow with time to greater than 1800 mg/l after 50 years. and the maximum transport of pollutants were about This means that the groundwater sustainable use at the 0.31 m/day. study area could be affected due to future increase of groundwater salinity.

Figure 14a: Calculated TDS concentration from MT3DMS model results with time.

Figure 14b: Calculated TDS concentration along El Mouhit drain route after 50 year.

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Results of MT3DMS model regarding nitrate be increased with time to greater than 80 mg/l after 50 groundwater (Figures 15a, b) indicated that the NO3 years. This means that NO3 concentration may violate concentration is about 80 mg/l in small reaches along the permissible limit of irrigation. This may affect and near the drain route, then decreases to 10 mg/l negatively sustainable use of groundwater in the study outside at a distance of 1 km far from the drain route. area. Predictions showed that the nitrate concentration could

Figure 15a: Calculated NO3 concentration from MT3DMS model results with time.

Figure 15b: Calculated NO3 concentration along El Mouhit drain route after 50 year.

7. Conclusions and recommendations between 633 mg/l and 1746 mg/l. Somewhat high The study area is located in the northwest of Giza concentrations of nitrate observed in drains ranging city. The main objective is to evaluate the groundwater from 48 mg/l to 88 mg/l referring to contamination quality status and the hazardous impacts for from agricultural and domestic wastewater discharged sustainable uses in the study area. into these drains. TDS in the groundwater samples The results indicated that TDS in drains ranges ranges from 612 mg/l to 4768 mg/l. The study area is

168 Nature and Science 2020;18(1) http://www.sciencepub.net/nature NSJ dominated by fresh to brackish groundwater, while Delta. Water and salt management in the Nile Delta: saline groundwater observed only in the southern and Report, (6). http://horizon.documentation.ird.fr/exl- southwestern parts. The groundwater is dominated by doc/pleins_textes/divers16-02/010066349.pdf. nitrate low concentrations (< 45 mg/l). High nitrate 3. APHA, 2017. Standard methods for the examination concentrations greater than 45 mg/l are found only in of water and wastewater, 23rd edition. Amer. Publ. the western and southwestern parts indicating Health Assoc., Amer. Water Works Assoc., Water contamination from domestic and agricultural Envir. Fed., AWWA catalog no: 10086, ISBN: wastewater in areas near of high vulnerability to 9780875532875. pollution. https://www.awwa.org/Store/Product- Details/productId/65266295. Visual MODFLOW simulation for groundwater 4. Balazov, A., Barokova, D., Mikulaz, K., Pfenderx, flow showed that the aquifer is recharged from excess D. and Soltesz, A. 2002. Numerical modelling of the irrigation water and leakage from irrigation network. groundwater flow in the left floodplain area of the MODPATH model indicated that the main Danube River. Proceedings of Algoritmy, 237-244. groundwater flow and also drain pollutants transport 5. Chao, D., Changlai, X., Xiujuan, L., Ji, L., Tonglin, from northeast to southwest and from east to north at X. and Guangjun, G. 2010. Numerical Simulation of wastewater treatment plant with a maximum velocity Groundwater Flow for Sustainable Utilization in Jixi of about 0.31 m/day. These indicate that the aquifer is City, China. IEEE, 978-1-4244-4713-8/10/ renewable and affected by surface activities. 6. EGPCO (The Egyptian General Petroleum MT3DMS model results regarding to TDS and Corporation), CONOCO (Conoco Coral), 1987. NO3 concentrations indicated increase of these Geological map of Egypt 1:500 000: NH 36 NW elements in groundwater with time. TDS concentration Cairo. Printed in Germany. is expected to increase to greater than 1800 mg/l after http://geospatial.com/products/series/geological- 50 years where the TDS of the groundwater was 612 scientific-maps/egypt-scale-1-500000-geological- maps-3000141/. ppm. Also, NO3 concentration is expected to increase to greater than 80 mg/l after 50 years. High 7. EGSA (Egyptian General Survey Authority), 1997. concentration occurred through the zone beneath the Topographic map of Egypt, Scale 1:50000”, Cairo drain pass and decreased outside confirming that west, NH 36-13a. 8. El-Araby, M., El Arabi, N., 2008. Modeling contaminants from agricultural and domestic wastes potential environmental impact of new settlements that migrate downward and may be extended into the on groundwater, Nile Delta, Egypt". unconfined portion of the aquifer system, which is 9. EMH (Egyptian Ministry of Health), 2007. high vulnerable to pollution. This means that the Ministerial decree on drinking water quality and the groundwater sustainable use could be affected by water quality for household use. Decree 458, May future quality changes. 2007. The following recommendations must be taken in http://documents.worldbank.org/curated/en/7022614 mind to avoid hazardous impacts of drainage water on 68233071240/pdf/E26430V30REVIS1IC10ES1ESI groundwater in the study area: AF1English.pdf.  It is utmost requirement for better 10. FAO, 1985.Water quality for agriculture. FAO management of wastewater and increasing the irrigation and drainage paper No. 29, Rev. 1, Rome, treatment degree to secondary or even tertiary degree. FAO.  Better management of using fertilizers in http://www.fao.org/docrep/003/t0234e/T0234E01.ht agriculture is very important. m#tab1.  Continuous monitoring for water quality 11. Farrag, K., Elbastamy, E., Ramadan, A., (2016) should be achieved. Health risk assessment of heavy metals in irrigated  Legislations should be acutely applied for agricultural crops, El-Saff Wastewater Canal, Egypt. conservation of water quality. Clean Soil Air Water 44(9):1085–1260.  Spreading public awareness through different 12. Freeze, R.A., Cherry, J.A., 1979. Groundwater. organization is important to minimize pollution. Prentice-Hall, Inc., Englewood Cliffs, U.S.A. 13. Khalaf, S., Gad, M.I., 2015. Modeling of

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